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Article

Bioaccumulation of Trace Elements in the Muscle of the Blackmouth Catshark Galeus melastomus from Mediterranean Waters

by
Samira Gallo
1,
Gianluca Nania
1,
Valentina Caruso
1,
Giorgia Zicarelli
2,
Francesco Luigi Leonetti
1,3,
Gianni Giglio
1,
Giorgio Fedele
1,
Chiara Romano
1,
Massimiliano Bottaro
3,
Olga Mangoni
4,
Danilo Scannella
5,
Sergio Vitale
5,
Fabio Falsone
5,
Giacomo Sardo
5,
Michele Luca Geraci
5,6,
Alessandra Neri
7,8,
Letizia Marsili
7,
Cecilia Mancusi
7,9,
Donatella Barca
1 and
Emilio Sperone
1,*
1
Department of Biology, Ecology and Earth Sciences, University of Calabria, Via P. Bucci, 87036 Rende, Italy
2
Department of Chemical, Biological, Pharmaceutical and Environmental Sciences, University of Messina, 98166 Messina, Italy
3
Department of Integrative Marine Ecology, Genoa Marine Centre, Anton Dohrn Zoological Station, 16126 Genoa, Italy
4
Department of Biology, University of Napoli Federico II, Complesso Universitario di Monte Sant’Angelo, 80134 Naples, Italy
5
Institute for Biological Resources and Marine Biotechnology (IRBIM), National Research Council CNR, Via Luigi Vaccara 61, 91026 Mazara del Vallo, Italy
6
Marine Biology and Fisheries Laboratory of Fano, Department of Biological, Geological and Environmental Sciences, University of Bologna, Viale Adriatico 1/n, 61032 Fano, Italy
7
Department of Environment, Earth and Physical Sciences, Siena University, Via Mattioli 4, 53100 Siena, Italy
8
Consorzio per il Centro Interuniversitario di Biologia Marina ed Ecologia Applicata “G. Bacci” (CIBM), Viale N. Sauro 4, 57128 Livorno, Italy
9
Environmental Protection Agency–Tuscany Region (ARPAT), Via Marradi 114, 57126 Livorno, Italy
*
Author to whom correspondence should be addressed.
Biology 2023, 12(7), 951; https://doi.org/10.3390/biology12070951
Submission received: 23 May 2023 / Revised: 28 June 2023 / Accepted: 30 June 2023 / Published: 3 July 2023
(This article belongs to the Special Issue Marine Wildlife and Biodiversity of the Mediterranean Sea: What's New?)
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Abstract

:

Simple Summary

This study examines the bioaccumulation of 17 trace elements (including aluminum, arsenic, cadmium, copper, and zinc, among others) in the muscle tissue of the blackmouth catshark (Galeus melastomus) from various locations in the Mediterranean Sea. This research focuses provides insights into the distribution and accumulation patterns of these elements in G. melastomus and sheds light on the potential risks posed by chemical contamination in the Mediterranean Sea. The study underscores the significance of investigating the impacts of pollutants on marine organisms, particularly sharks, to develop effective conservation and management strategies. The data contribute to our understanding of trace element bioaccumulation in elasmobranch species, thus highlighting the importance of protecting these key ecological players in marine ecosystems.

Abstract

Environmental pollution, particularly in the marine environment, has become a significant concern due to the increasing presence of pollutants and their adverse effects on ecosystems and human health. This study focuses on the bioaccumulation of trace elements in the muscle tissue of the blackmouth catshark (Galeus melastomus) from different areas in the Mediterranean Sea. Trace elements are of interest due to their persistence, toxicity, and potential for bioaccumulation. This research aims to assess the distribution and accumulation of trace elements in the muscle tissue of G. melastomus and investigate their potential impact on the deep-sea environment of the Mediterranean. The focused areas include the Ligurian Sea, the northern and central Tyrrhenian Sea, the southern Tyrrhenian Sea, the Ionian Sea, the Pantelleria Waters, and the Gela Waters. Samples were collected following established protocols, and trace element analysis was conducted using inductively coupled plasma mass spectrometry. The study provides data on the concentrations of 17 trace elements, namely aluminum, arsenic, cadmium, cobalt, copper, manganese, molybdenum, nickel, zinc, selenium, strontium, lead, chromium, iron, barium, bismuth, and uranium. The findings contribute to a better understanding of trace element bioaccumulation patterns in elasmobranch species, specifically G. melastomus, and highlight the potential risks associated with chemical contamination in the Mediterranean Sea. This research emphasizes the importance of studying the impacts of pollutants on marine organisms, particularly those occupying key ecological roles, like sharks, to support effective conservation and management strategies.

1. Introduction

Environmental pollution is an issue of particular interest to the scientific community due to the drastic increase of pollutants in the environment observed in the last decade [1]. Pollution in the marine environment is a global concern owing to the devastating effects of contaminants, which are bioaccumulated and sometimes biomagnified through trophic webs up to humans [2]. Biomagnification results in the dispersal of pollutants far from their point of origin and areas affected by intense human activities (e.g., [3,4,5]).
Trace elements are frequently assessed due to their high persistence, toxicity, and bioaccumulation affinities [6]. The World Health Organization (WHO) has divided these compounds into essential and non-essential categories: while the former play a fundamental role in biological systems (i.e., I, Zn, Se, Fe, Cu, Cr, and Mo) and could become toxic beyond a certain threshold [7], the latter do not play any physiological roles and are often toxic even at low concentrations (i.e., Hg, Pb, and Cd) [8]. Other elements (e.g., Mn, Co, As, Ni, or V) are defined by some authors as potentially essential [9].
Trace elements adsorbed onto aeolian particles and river particulates [10] are capable of being transported over long distances [11,12], and upon contact with the sea surface, some can dissolve in the upper water masses [13]. In addition, a trace element fraction, through biological processes, may reach the ocean floor as particulate matter, where they can be incorporated into sediments [14,15]. Among trace element sources in the Mediterranean Sea, aerosol powders [16] and river particulates [10] have been identified in the first 100 m of waters columns and in deep deposits (300–600 m) [14]
The tissue accumulation of trace elements depends on an organism’s water uptake. It can occur either via direct contact (e.g., through the epidermis, gills, and digestive tract) or diet [17]. Several factors influence element accumulation, such as uptake pathways, tissue function, physiological exposure, reproductive activity, life stage, and sex [18,19,20,21]; thus, this process is highly variable. Trace elements and metals that cannot be excreted are retained in the body, where they are perpetually added to over the life span of the organism [22,23]. Since marine organisms are able to accumulate trace elements, they are often considered relatively good semi-quantitative bioindicators, reflecting the occurrence and bioavailability of contaminants in the areas where they live [24].
Sharks are mostly long-lived elasmobranch species and occupy apex–meso-predator roles in their respective food webs (e.g., [25]). Therefore, they are known to accumulate high levels of metals, metalloids, and other pollutants in their tissues [26,27,28]. This feature results in deleterious effects on their normal physiology/biochemistry (e.g., immune and endocrine toxicity, reproductive deficits and tumor promotion) and ultimately on shark population dynamics [29,30,31]. Given their key role in aquatic ecosystems, especially in a closed basin such as the Mediterranean, it is crucial to study how contaminants affect these organisms [1,32].
Available information regarding the bioaccumulation of pollutants in elasmobranchs is currently limited to either specific locations of the world or to a restricted number of species [26,33,34]. Despite sharks are not being considered a popular source of fish meat [35], several shark species are targeted by fisheries to satisfy market demands for food consumption [36,37], thus raising public health concerns about the chemical contamination in elasmobranch tissues [38,39]. In particular, elasmobranchs in the Mediterranean Sea have mostly been considered low-economic bycatches and even a nuisance in the past and thus massively discarded, as in the case of the Galeus melastomus (Rafinesque, 1810) in the South of Sicily [40,41,42]. This small-sized shark lives in deep waters from 150 to more than 2000 m [43,44], even though it can be occasionally (especially juveniles) found over the inner shelf (50–60 m) [37,43,45,46]. G. melastomus feeds mainly on shelf-living species and natantian and reptantian crustaceans, as well as with teleosts and occasionally galley leftovers [47] and even birds [48]. Given the important role of the elasmobranchs in the marine ecosystem equilibrium and the paucity of data, the aim of this paper is to fill a knowledge gap by investigating and comparing the accumulation of trace elements pollutants in the muscle of the blackmouth catshark from seven areas in the Mediterranean Sea. This will contribute to assessing a potential benchmark to evaluate the impact of these elements on the Mediterranean deep-sea environment.

2. Materials and Methods

2.1. Catshark Batch and Sampling Methodology

The study area is the western–central Mediterranean Sea, which includes the northern Tyrrhenian and Ligurian Sea (geographical sub-area, GSA 9), the central and southern Tyrrhenian Sea (GSA 10), the Ionian Sea (GSA 19), and the South of Sicily (GSA 16) (Figure 1). The northern part of the Tyrrhenian Sea (GSA 9) is more heterogeneous from a ecological and morphological point of view, and the continental shelf extends up to 150 m and to a maximum depth of between 2000 and 2200 m. The southern–central Tyrrhenian Sea (GSA 10) is characterized by two principal abyssal plains with a maximum depth between 2900 and 3600 m and by the presence of two important submarine volcanos. The principal currents in the GSA 9 originate from the wind, and they are subjected to significant seasonal variations, while the geophysical, morphological, and dynamic structures of the GSA 10 are one of the most complex of all the Italian peninsulas [49,50]. The Ionian Sea (GSA 19) is the deepest sea of the entire Mediterranean Basin with a mean depth of ca. 2000 m. The Taranto Valley divides the Ionian Sea into the western and the south-eastern slopes [51] The Strait of Messina marks the boundary between the Tyrrhenian and the Ionian Seas, where strong vertical gradients, horizontal gradients, and tidal currents originate [52]. The Strait of Sicily (GSA 16) is an area of transition between the sub-basins of the western and eastern Mediterranean and includes the Sicilian and Tunisian platforms. The geomorphology is very complex, characterized by several sea mountains (banks) composed of sedimentary or volcanic rocks, such as the volcanic island of Pantelleria located between the Sicilian and Tunisian platforms. This topography affects the currents around the banks, resulting in significant upwelling, which, in turn, increases overall productivity, making this channel one of the most important biodiversity hotspots in the Mediterranean basin [53].
The specimens of the GSA9 and GSA16 were collected during the international bottom trawl survey in the Mediterranean (MEDITS), while the samples of the GSA10 and GSA19 were collected via commercial bottom trawling. In Table 1, geographical coordinates, sampling period, number of specimens, and catching depth are reported. Specimens of G. melastomus were collected following the Italian law “Decreto Legislativo 4 marzo 2014, n. 26”, which implemented the “European Directive 2010/63/UE” and is recognized as using the guidelines put forward in Ebert et al. [54].

2.2. Tissue Dissection

The specimens—previously stored at −20 °C—were thawed at room temperature for 24 h prior for further manipulation [55]. Each sample was photographed, and its sex and biometric measurements were recorded: fresh weight (W), total length (TL), and fork length (FL). W was taken to the nearest 0.01 g whereas TL to the 0.1 cm. Subsequently, the specimens were dissected using surgical stainless steel straight scissors with alternating tips, precision stainless steel tweezers, and disposable surgical scalpels (measures n.10 and n.11). A cut was made ventrally, from the cloacal opening up to the cardiac cavity. Muscle biopsies were taken from both sides, below the peritoneal membrane, up to about 1 gr each side, and the samples were stored in dry conditions (−20 °C) in 1.5 mL Eppendorf tubes until analysis.

2.3. Analysis of Trace Elements

The analysis provided the concentrations, expressed in ppb (parts per billion), of 17 trace elements: aluminum (Al), arsenic (As), cadmium (Cd), cobalt (Co), copper (Cu), manganese (Mn), molybdenum (Mo), nickel (Ni), zinc (Zn), selenium (Se), strontium (Sr), lead (Pb), chromium (Cr), iron (Fe), barium (Ba), bismuth (Bi), and uranium (U). This analysis was conducted using an inductively coupled plasma mass spectrometer (ICP-MS, PerkinElmer, ElanDRCe model). The DRC consists of a quadrupole placed inside an enclosed reaction chamber. This quadrupole eliminates polyatomic interferences caused by the combination of plasma gases and sample matrix constituents before they can enter the analyzing quadrupole. This ion-molecule chemistry uses a reaction gas (CH4) to “chemically scrub” polyatomic or isobaric species from the ion beam before they enter the analyzer, resulting in improved detection limits for traditionally difficult elements, including As, Cr, Fe, Se, and others. The plasma torch, however, is powered using Argon with a purity of 5.00. The strength of this equipment is its fast multiplexing, allowing the acquisition of the data of several elements at once with high precision.
Prior to analysis, in order to solubilize the samples, muscle tissue samples were chemically digested, according to the protocol of De Donato et al. [56], and is described as follows: (a) Drying—the tissue was air dried in a laminar flow hood (Herasafe, model KS-12 class II) for 24 h. (b) Weighing—each sample was weighed in its Teflon (TFM) digestion vessel on an analytical balance with the sensitivity of 0.0001 (g) (Sartorius, model CP324S-0CE). (c) Acid digestion—12 mL of ultrapure HNO3 (64–69%) was added to the tissue, the vessels (hermetically sealed) were installed on a carousel and placed inside an EMC microwave oven (Mars 6). A program that provides a rising temperature ramp up to 180 °C was then applied for 20 min, followed by 20 min of cooling. After cooling, the vessels were worn out. (d) Evaporation—the content was transferred from the digestion vessel into larger vessels, taking care to rinse any residue with ultra-pure water (UPW). These vessels were then placed on a hot plate at 200 °C for about 2–3 h (t changes according to the starting volume) in order to eliminate acid fumes and to avoid damage to the instrumentation used for analysis. (e) Make up to the mark—the concentrated solution obtained by evaporation was transferred into glass matrasses and diluted to the volume of 100 mL using ultra-pure water. The solution was then homogenized inside the matrasses by shaking (manual stirring) in order to avoid the uneven distribution of the elements at the bottom of the flask. (f) Storage—the solution was temporarily stored in sterile containers at 4 °C until analysis.
During phases (a) and (b), the muscles’ water percentage was also measured, thus allowing the conversion of the dry weight values, returned by the ICP-MS, to wet weight (mg/Kg), using the equation of Gaion et al. [57]:
WW = DW × (1 − WP)
where WW is the wet weight, DW is the dry weight, and WP is the water percentage loss during the drying stage. The blank was prepared with ultra-pure water and ultrapure nitric acid (100 µL HNO3:10 mL UPW). The internal standard (Re) was added to both blank, standard, and other solutions. The ICP-MS was calibrated using the ICP multi-element standard solution VI for ICP-MS (Merck). The accuracy of the method was evaluated using the Lobster Hepatopancreas (Tort-3; National Research Council Canada) as the certified reference material (CRM). The same preparation procedure was used on the CRM and these solutions were used as unknown samples during the analytical sequence. During the analysis, the blank and the CRM were processed by the ICP-MS at the beginning and at the end and were also interspersed with every six samples (checking that the values were always in the norm and that the drift of the instrument did not affect the results obtained). Accuracies were better than 8%, with most elements within ±5%. The detection limit was set at three times the standard deviation of the blanks and its value oscillated around 0.2 mg/Kg.

2.4. Data Analysis

For the comparison of trace elements mean values between sexes and among areas, the Mann–Whitney U-test and Kruskal–Wallis test were used, respectively, with Dunn test as the post hoc test. To investigate a possible correlation between trace element concentration and the growth of the species, the bioaccumulation of each area was compared to the TL of the specimens by means of linear regression. All statistical analyses were carried out using the Instat 3.0 program. We considered five significance levels: no significance (NS, p > 0.05), not quite significant (§, 0.05 ≤ p ≤ 0.01), significant (*, 0.01 ≤ p ≤ 0.001), very significant (**, 0.001 ≤ p < 0.0001), and extremely significant (***, p ≤ 0.0001). In addition, the trace element pollution index (TEPI) was calculated as stated by Richir and Gobert [58]:
TEPI = (Cf1 × Cf2 … Cfn)1/n
where Cfn is the normalized mean concentration of the trace element—calculated as the mean concentration of each TE per location divided by the overall mean of that TE—and n is the total number of examined potentially toxic elements [59]. Once the TEPI values have been calculated, they can be classified qualitatively according to a three-level contamination scale, defined by the quartile method [59].

3. Results

The batch of samples was composed of 78 specimens with a total of 38 females and 40 males, including 68 animals in the adult size class (TL > 34 cm) and 10 in the sub-adult size class (23 cm > TL > 34 cm), according to Ebert et al. [54]. The mean values of TL, W, and sample size are reported in Table 2.
The results obtained for 17 trace elements were grouped by sex and areas. The average values of DW concentrations (mg/Kg) were summarized in Table 3.
On the basis of the average concentration values per element, males tended to show higher values than females; however, the Mann–Whitney U-test shows a statistically significant difference only for As (*, p < 0.01) (Figure 2). The specimens originating from the CT and the LS showed greater bioaccumulation—six elements each—while the specimens from PW showed higher bioaccumulation values of Al. The samples originating from GW waters showed the lowest bioaccumulation—12 elements. In more detail, Figure 3 highlights the number of elements of which the different areas showed higher concentrations when compared to the other sites.
As for the comparison of the trace elements between different areas (Table 4), specimens from the Pantelleria Waters (PW) showed a statistically significant difference in five of the elements (Al, As, Cd, Co, and Pb; p < 0.0001), while the specimens from Gela Waters (GW) showed a statistically significant difference in six elements (As, Cd, Co, Cu, Pb, and Zn; p < 0.0001). Moving to the Tyrrhenian Sea areas (GSA 9 and 10), specimens from ST showed no statistically significant differences, whereas those caught in CT, NT, and LS areas displayed statistically significant differences in five (Al, Fe, Mn, Se, and Sr; 0.03 < p < 0.0001), three (Bi, Sr, and U; p < 0.0001), and six (Al, Cr, Mo, Ni, Se and Sr; 0.02 < p < 0.0001) elements, respectively. Finally, the specimens originating from the GSA 19 (IS) differed in two elements (Ba, p < 0.0001, and Fe, p < 0.03).
Regarding the relationship between trace elements and the growth of the species, As was the only significant element in every area, with a positive trend (i.e., the concentrations for this element increases with increasing TL), while five elements (Cd, Cr, Cu, Mo, and Zn) showed a negative trend or no trends across all sites. Specimens from CT showed the greatest statistical significance—in nine elements—and the greatest number of negative trends. In general, despite slight differences between areas, more negative correlations were observed. Statistical results are summarized in Figure 4.
Scales of abundance for each sex, sampling areas, and overall amounts (Table 5) are obtained using concentration mean values.
Taking into account the most abundant elements found (As, Fe, Al, Zn, Sr, Cr, Cu, Mn, and Ni) and the two elements within the Regulations EC No 1881/2006 (Cd and Pb), we calculated the mean concentrations for the WW and determined the percentages of contribution for each area (Figure 5). The 100% refers to the total amount of each element obtained, so that the concentration per site can be observed in percentage and the comparison between locations is visible.
The water percentage in muscles was found to be 70.45% (average), then the average values of the concentrations for the WW were obtained.
TEPI was calculated and reported in Figure 6. The first and third quartiles were used as thresholds to classify the level of contamination impact and they were equal to 0.563 and 0.997, respectively. The sites PW and GW were found to be the least affected by trace element pollution (TEPI < first quartile) while the sites CT and LS were the most impacted (TEPI > third quartile). The areas ST, IS, NT, and LS stood in the middle of the contamination scale (first quartile > TEPI< third quartile).

4. Discussion

Although previous studies on bioaccumulation for G. melastomus in the Mediterranean Sea are indeed present in the literature, e.g., [57,60,61], our study is, to the best of our knowledge, the first to have compared many trace elements (17) across different sites (7).
Males showed a trend for higher mean values for the concentration of trace elements than females, supporting previously published findings that described a lower bioaccumulation in females of many species.
Energy investment during reproduction, the size at which they reach sexual maturity, the energy cost of gamete synthesis, and the transfer of contaminants during oocyte development, have all been suggested as putative explanations for the observed sexual dimorphic variation [57,62].
Interestingly, females showed a very high bioaccumulation of As, which is one of the most controversial elements. According to the WHO, As is classified as potentially essential. Its presence in the water can originate from both natural and anthropogenic sources, and numerous studies investigating human toxicity are underway. Storelli et al. [63] had already reported a positive correlation between body size and the bioaccumulation of As, further confirmed by our results.
Both sexes showed an identical bioaccumulation of Pb with no significant differences. This non-essential element can be toxic to marine organisms as well as humans, even at low concentrations [8]. The accumulation begins at the embryonic stage [64]—if the egg is exposed to this pollutant—and it continues through subsequent developmental stages via ingestion (mainly through prey [65]). However, it is an elements that can be expelled from the body throughout an animal’s life [66,67].
In terms of areas, CT and LS specimens showed the highest bioaccumulation (35.3% each), followed by IS specimens, then NT, ST and finally PW. These differences could be explained by the hydrodynamic conditions that characterize the various areas, as observed in other contexts [68,69]. Nevertheless, the excellent difference in bioaccumulation rates in PW and GW compared to all the other areas stands out in particular. Two reasons could be proposed to justify this result. First of all, both large and mesoscale oceanographic patterns in the Sicilian Channel are strongly related to the combining effects of wind and seafloor topography; in particular, wind-induced coastal upwelling along the southern Sicilian coast could impact the pollution dispersion toward the east [70,71,72]. The removal of pollutants towards the east could therefore limit their bioaccumulation, especially in demersal species. Secondly, they could simply be more remote areas and therefore subject to low levels of pollution.
The correlation between trace elements and growth has showed an overall negative trend, probably due to a change in diet (in cases where food was the main source), a possible “moving away” dispersal from the source or to the mechanisms of metabolization and the expulsion of pollutants that developed during growth (e.g., development of oocytes and deposition). It is worth noting that while samples from most sites do not have a wide variety of lengths (TL > 34 cm), only the central Tyrrhenian Sea batch included sub-adults (23.6 < TL < 51.0 cm). The results of the present study showed values for Cd and Pb equal to 0.023 mg/Kg (WW) and 0.029 mg/Kg (WW), respectively. Both values exhibited below maximum levels for certain contaminants in foodstuffs (Cdlimit = 0.050 mg/Kg; Pblimit = 0.30 mg/Kg) set by the “Commission Regulation (EC) No 1881/2006 of 19th December 2006”, suggesting that the levels of this trace element in blackmouth catshark in the western–central Mediterranean Sea are safe for human consumption.
By comparing the As content in the blackmouth catshark with previous studies, we found that the mean value at our sites (2020–2021) is 27.004 mg/Kg WW (91.383 mg/Kg DW), as opposed to the quantified maximum value in the Aegean Sea of 13.07 mg/Kg WW reported in Storelli and Marcotrigiano [60] in other Mediterranean areas (two in the Adriatic Sea, one in the Ionian Sea, and one in the Aegean Sea).
Focusing only on the northern Tyrrhenian Sea, the elements As, Cd, Pb, and Cu appeared in amounts of 121.07 mg/Kg, 0.14 mg/Kg, 0.16 mg/Kg, and 1.75 mg/Kg, respectively. Previously, Gaion et al. [57] found greater values for As and Pb (174.5 mg/Kg and 0.35 mg/Kg) and almost equal or slightly lower values for Cd and Cu (0.1 mg/Kg and 1.7 mg/Kg).
Mille et al. [61] analyzed two different populations of G. melastomus—one in the Mediterranean Sea (Gulf of Lions) and one in the Atlantic Ocean (Bay of Biscay). The comparison between the mean values of their populations (Atlantic and Mediterranean) and our seven areas from the western–central Mediterranean Sea showed higher concentrations for the specimens of the present study, i.e., Cd, Pb, Zn, and Ni, while the average of our values for Cu was lower than the average they obtained in the Mediterranean Sea.
Furthermore, the trace elements pollution index (TEPI) for the western–central Mediterranean Sea (0.873) estimated in the present study yielded results that were lower than those reported by Mille et al. [61] in the northern–western Mediterranean Sea (1.13). Instead, the lower values obtained in the GSA 16 (PW = 0.563 and GW = 0.488) were similar to those observed in the northern–eastern Atlantic Ocean (0.7) and in the Bay of Biscay (0.56).

5. Conclusions

In conclusion, these results enrich our knowledge about this deep-water species and provide more insights into the condition of the Mediterranean Sea’s environment in terms of pollution by trace elements. This study, nevertheless, represents a starting point for further studies, aimed at deepening our understanding of what occurs in different tissues and what the consequences for human health could be.

Author Contributions

Conceptualization, E.S., D.B., L.M., C.M., O.M., M.B. and M.L.G.; methodology, D.B., E.S., M.B., O.M., C.M. and M.L.G.; formal analysis, S.G., G.G., G.F., M.L.G. and S.V.; investigation, S.G., G.N., V.C., G.Z., F.L.L., C.R., D.S., S.V., F.F., G.S., A.N. and C.M.; resources, M.B., D.B., S.V. and E.S.; data curation, S.G., G.Z., C.R., G.G., G.F., M.L.G., A.N. and C.M.; writing—original draft preparation, S.G., G.N., V.C., C.M., D.B. and E.S.; writing—review and editing, G.F., F.L.L., M.B., O.M., D.S., S.V., F.F., G.S. and M.L.G.; supervision, E.S., D.B., M.B., O.M. and L.M.; funding acquisition, M.B., E.S. and D.B. All authors have read and agreed to the published version of the manuscript.

Funding

This research was funded by Stazione Zoologica “A. Dohrn”, in the ambit of the CRIMAC project “SECRETS from CALABRIA”.

Institutional Review Board Statement

The chondrichthyan specimens enrolled in the present work were obtained from commercial fisheries. The activity was conducted under the conditions of the Regulation of the European Parliament and the Council for fishing in the General Fisheries Commission for the Mediterranean (GFCM) Agreement area and amended Council Regulation (EC) No. 1967/2006. All procedures were carried out with the approval of the “Ministero della transizione ecologica—MiTE” (n. authorization 0008263, 25 January 2022).

Informed Consent Statement

Not applicable.

Data Availability Statement

Data are available on request due to restrictions, e.g., privacy or ethical.

Acknowledgments

The authors are grateful to the professional fishermen who provided specimens and to Luigi Passarelli, Pina Lucia Cacciola, and Victor Pepe Bellomo for their help during collection and analysis.

Conflicts of Interest

The authors declare no conflict of interest.

References

  1. Consales, G.; Marsili, L. Assessment of the Conservation Status of Chondrichthyans: Underestimation of the Pollution Threat. Eur. Zool. J. 2021, 88, 165–180. [Google Scholar] [CrossRef]
  2. Landrigan, P.J.; Stegeman, J.J.; Fleming, L.E.; Allemand, D.; Anderson, D.M.; Backer, L.C.; Brucker-Davis, F.; Chevalier, N.; Corra, L.; Czerucka, D.; et al. Human Health and Ocean Pollution. Ann. Glob. Health 2020, 86, 151. [Google Scholar] [CrossRef]
  3. Holsbeek, L.; Joiris, C.R.; Debacker, V.; Ali, I.B.; Roose, P.; Nellissen, J.P.; Gobert, S.; Bouquegneau, J.M.; Bossicart, M. Heavy Metals, Organochlorines and Polycyclic Aromatic Hydrocarbons in Sperm Whales Stranded in the Southern North Sea During the 1994/1995 Winter. Mar. Pollut. Bull. 1999, 38, 304–313. [Google Scholar] [CrossRef]
  4. Solé, M.; Porte, C.; Albaigés, J. Hydrocarbons, PCBs and DDT in the NW Mediterranean Deep-Sea Fish Mora Moro. Deep. Sea Res. Part I Oceanogr. Res. Pap. 2001, 48, 495–513. [Google Scholar] [CrossRef]
  5. Kucklick, J.R.; Struntz, W.D.J.; Becker, P.R.; York, G.W.; O’Hara, T.M.; Bohonowych, J.E. Persistent Organochlorine Pollutants in Ringed Seals and Polar Bears Collected from Northern Alaska. Sci. Total Environ. 2002, 287, 45–59. [Google Scholar] [CrossRef]
  6. Naser, H.A. Assessment and Management of Heavy Metal Pollution in the Marine Environment of the Arabian Gulf: A Review. Mar. Pollut. Bull. 2013, 72, 6–13. [Google Scholar] [CrossRef]
  7. Amiard, J.C.; Pineau, A.; Boiteau, H.L.; Metayer, C.; Amiard-Triquet, C. Application de La Spectrometrie d’absorption Atomique Zeeman Aux Dosages de Huit Elements Traces (Ag, Cd, Cr, Cu, Mn, Ni, Pb et Se) Dans Des Matrices Biologiques Solides. Water Res. 1987, 21, 693–697. [Google Scholar] [CrossRef]
  8. Nordberg, G.F. Historical Perspectives on Cadmium Toxicology. Toxicol. Appl. Pharm. 2009, 238, 192–200. [Google Scholar] [CrossRef] [PubMed]
  9. Guéguen, M.; Amiard, J.C.; Arnich, N.; Badot, P.M.; Claisse, D.; Guérin, T.; Vernoux, J.P. Shellfish and Residual Chemical Contaminants: Hazards, Monitoring, and Health Risk Assessment along French Coasts. Rev. Environ. Contam. Toxicol. 2011, 213, 55–111. [Google Scholar] [CrossRef]
  10. Martin, J.M.; Elbaz-Poulichet, F.; Guieu, C.; Loÿe-Pilot, M.D.; Han, G. River versus Atmospheric Input of Material to the Mediterranean Sea: An Overview. Mar. Chem. 1989, 28, 159–182. [Google Scholar] [CrossRef]
  11. Nriagu, J.O. Natural Sources of Trace Metals in the Atmosphere: Global Assessment. Nature 1989, 338, 47–49. [Google Scholar] [CrossRef]
  12. Buat-Ménard, P. Global Change in Atmospheric Metal Cycles. In Global Atmospheric Chemical Change; Springer: Dordrecht, The Netherlands, 1993; pp. 271–311. [Google Scholar] [CrossRef]
  13. Flegal, A.R.; Patterson, C.C. Vertical Concentration Profiles of Lead in the Central Pacific at 15°N and 20°S. Earth Planet. Sci. Lett. 1983, 64, 19–32. [Google Scholar] [CrossRef]
  14. Veron, A.; Lambert, C.E.; Isley, A.; Linet, P.; Grousset, F. Evidence of Recent Lead Pollution in Deep North-East Atlantic Sediments. Nature 1987, 326, 278–281. [Google Scholar] [CrossRef]
  15. Hamelin, B.; Grousset, F.E.; Biscaye, P.E.; Zindler, A.; Prospero, J.M. Lead Isotopes in Trade Wind Aerosols at Barbados: The Influence of European Emissions over the North Atlantic. J. Geophys. Res. Ocean. 1989, 94, 16243–16250. [Google Scholar] [CrossRef]
  16. Bard, E.; Hamelin, B.; Fairbanks, R.G.; Zindler, A. Calibration of the 14C Timescale over the Past 30,000 Years Using Mass Spectrometric U–Th Ages from Barbados Corals. Nature 1990, 345, 405–410. [Google Scholar] [CrossRef] [Green Version]
  17. Mathews, T.; Fisher, N.S. Dominance of Dietary Intake of Metals in Marine Elasmobranch and Teleost Fish. Sci. Total Environ. 2009, 407, 5156–5161. [Google Scholar] [CrossRef]
  18. Le Croizier, G.; Schaal, G.; Gallon, R.; Fall, M.; Le Grand, F.; Munaron, J.M.; Rouget, M.L.; Machu, E.; Le Loc’h, F.; Laë, R.; et al. Trophic Ecology Influence on Metal Bioaccumulation in Marine Fish: Inference from Stable Isotope and Fatty Acid Analyses. Sci. Total Environ. 2016, 573, 83–95. [Google Scholar] [CrossRef] [Green Version]
  19. Anandkumar, A.; Nagarajan, R.; Prabakaran, K.; Bing, C.H.; Rajaram, R. Human Health Risk Assessment and Bioaccumulation of Trace Metals in Fish Species Collected from the Miri Coast, Sarawak, Borneo. Mar. Pollut. Bull. 2018, 133, 655–663. [Google Scholar] [CrossRef]
  20. Annabi, A.; El Mouadeb, R.; Herrel, A. Distinctive Accumulation Patterns of Heavy Metals in Sardinella Aurita (Clupeidae) and Mugil Cephalus (Mugilidae) Tissues. Environ. Sci. Pollut. Res. Int. 2018, 25, 2623–2629. [Google Scholar] [CrossRef]
  21. Kalantzi, I.; Mylona, K.; Pergantis, S.A.; Coli, A.; Panopoulos, S.; Tsapakis, M. Elemental Distribution in the Different Tissues of Brood Stock from Greek Hatcheries. Aquaculture 2019, 503, 175–185. [Google Scholar] [CrossRef]
  22. Gray, J.S. Biomagnification in Marine Systems: The Perspective of an Ecologist. Mar. Pollut. Bull. 2002, 45, 46–52. [Google Scholar] [CrossRef]
  23. Wang, W.X. Interactions of Trace Metals and Different Marine Food Chains. Mar. Ecol. Prog. Ser. 2002, 243, 295–309. [Google Scholar] [CrossRef] [Green Version]
  24. Raknuzzaman, M.; Ahmed, M.K.; Islam, M.S.; Habibullah-Al-Mamun, M.; Tokumura, M.; Sekine, M.; Masunaga, S. Trace Metal Contamination in Commercial Fish and Crustaceans Collected from Coastal Area of Bangladesh and Health Risk Assessment. Environ. Sci. Pollut. Res. 2016, 23, 17298–17310. [Google Scholar] [CrossRef] [PubMed]
  25. Heupel, M.R.; Knip, D.M.; Simpfendorfer, C.A.; Dulvy, N.K. Sizing up the Ecological Role of Sharks as Predators. Mar. Ecol. Prog. Ser. 2014, 495, 291–298. [Google Scholar] [CrossRef] [Green Version]
  26. Giovos, I.; Brundo, M.V.; Doumpas, N.; Kazlari, Z.; Loukovitis, D.; Moutopoulos, D.K.; Spyridopoulou, R.N.A.; Papadopoulou, A.; Papapetrou, M.; Tiralongo, F.; et al. Trace Elements in Edible Tissues of Elasmobranchs from the North Aegean Sea (Eastern Mediterranean) and Potential Risks from Consumption. Mar. Pollut. Bull. 2022, 184, 114129. [Google Scholar] [CrossRef]
  27. Reinero, F.R.; Milazzo, C.; Minervino, M.; Marchio, C.; Filice, M.; Bevacqua, L.; Giglio, G.; Leonetti, F.L.; Micarelli, P.; Tripepi, S.; et al. Parasitic Load, Hematological Parameters, and Trace Elements Accumulation in the Lesser Spotted Dogfish Scyliorhinus Canicula from the Central Tyrrhenian Sea. Biology 2022, 11, 663. [Google Scholar] [CrossRef]
  28. Reinero, F.R.; Becerril-Garcìa, E.E.; Elorriagaverplancken, F.R.; Melo-Barrera, F.N.; Toraldo-Serra, M.L.; Giglio, G.; Micarelli, P.; Tripepi, S.; Galvan-Magana, F.; Sperone, E. Stable Isotopes Provide Evidence of a Trophic Shift in the Lesser Spotted Dogfish Scyliorhinus Canicula from the Central Tyrrhenian Sea. Mediterr. Mar. Sci. 2023, 24, 1–6. [Google Scholar] [CrossRef]
  29. Storelli, M.M.; Barone, G.; Santamaria, N.; Marcotrigiano, G.O. Residue Levels of DDTs and Toxic Evaluation of Polychlorinated Biphenyls (PCBs) in Scyliorhinus Canicula Liver from the Mediterranean Sea (Italy). Mar. Pollut. Bull. 2006, 52, 696–700. [Google Scholar] [CrossRef] [PubMed]
  30. Alves, L.M.F.; Nunes, M.; Marchand, P.; Le Bizec, B.; Mendes, S.; Correia, J.P.S.; Lemos, M.F.L.; Novais, S.C. Blue Sharks (Prionace Glauca) as Bioindicators of Pollution and Health in the Atlantic Ocean: Contamination Levels and Biochemical Stress Responses. Sci. Total Environ. 2016, 563–564, 282–292. [Google Scholar] [CrossRef]
  31. Filice, M.; Reinero, F.R.; Cerra, M.C.; Faggio, C.; Leonetti, F.L.; Micarelli, P.; Giglio, G.; Sperone, E.; Barca, D.; Imbrogno, S. Contamination by Trace Elements and Oxidative Stress in the Skeletal Muscle of Scyliorhinus Canicula from the Central Tyrrhenian Sea. Antioxidants 2023, 12, 524. [Google Scholar] [CrossRef]
  32. Bevacqua, L.; Reinero, F.R.; Becerril-García, E.E.; Elorriaga-Verplancken, F.R.; Juaristi-Videgaray, D.; Micarelli, P.; Galván-Magaña, F.; Curiel-Godoy, P.; Giglio, G.; Tripepi, S.; et al. Trace Elements and Isotopes Analyses on Historical Samples of White Sharks from the Mediterranean Sea. Eur. Zool. J. 2021, 88, 132–141. [Google Scholar] [CrossRef]
  33. Cullen, J.A.; Marshall, C.D.; Hala, D. Integration of Multi-Tissue PAH and PCB Burdens with Biomarker Activity in Three Coastal Shark Species from the Northwestern Gulf of Mexico. Sci. Total Environ. 2019, 650, 1158–1172. [Google Scholar] [CrossRef]
  34. Boldrocchi, G.; Monticelli, D.; Omar, Y.M.; Bettinetti, R. Trace Elements and POPs in Two Commercial Shark Species from Djibouti: Implications for Human Exposure. Sci. Total Environ. 2019, 669, 637–648. [Google Scholar] [CrossRef]
  35. Almeida, C.; Karadzic, V.; Vaz, S. The Seafood Market in Portugal: Driving Forces and Consequences. Mar. Policy 2015, 61, 87–94. [Google Scholar] [CrossRef] [Green Version]
  36. Falsone, F.; Scannella, D.; Geraci, M.L.; Vitale, S.; Colloca, F.; Di Maio, F.; Milisenda, G.; Gancitano, V.; Bono, G.; Fiorentino, F. Identification and Characterization of Trammel Net Métiers: A Case Study from the Southwestern Sicily (Central Mediterranean). Reg. Stud. Mar. Sci. 2020, 39, 101419. [Google Scholar] [CrossRef]
  37. Bradai, M.N.; Saidi, B.; Enajjar, S. Overview on Mediterranean Shark’s Fisheries: Impact on the Biodiversity. In Marine Ecology—Biotic and Abiotic Interactions; IntechOpen: London, UK, 2018. [Google Scholar] [CrossRef] [Green Version]
  38. Mull, C.G.; Lyons, K.; Blasius, M.E.; Winkler, C.; O’Sullivan, J.B.; Lowe, C.G. Evidence of Maternal Offloading of Organic Contaminants in White Sharks (Carcharodon Carcharias). PLoS ONE 2013, 8, e62886. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  39. Sumpter, J.P. Protecting Aquatic Organisms from Chemicals: The Harsh Realities. Philos. Trans. A Math. Phys. Eng. Sci. 2009, 367, 3877–3894. [Google Scholar] [CrossRef]
  40. Ragonese, S.; Vitale, S.; Dimech, M.; Mazzola, S. Abundances of Demersal Sharks and Chimaera from 1994-2009 Scientific Surveys in the Central Mediterranean Sea. PLoS ONE 2013, 8, e74865. [Google Scholar] [CrossRef] [Green Version]
  41. Geraci, M.L.; Ragonese, S.; Norrito, G.; Scannella, D.; Falsone, F.; Vitale, S. A Tale on the Demersal and Bottom Dwelling Chondrichthyes in the South of Sicily through 20 Years of Scientific Survey. In Chondrichthyes—Multidisciplinary Approach; InTech: London, UK, 2017. [Google Scholar]
  42. Falsone, F.; Gancitano, V.; Geraci, M.L.; Sardo, G.; Scannella, D.; Serena, F.; Vitale, S.; Fiorentino, F. Assessing the Stock Dynamics of Elasmobranchii off the Southern Coast of Sicily by Using Trawl Survey Data. Fishes 2022, 7, 136. [Google Scholar] [CrossRef]
  43. Ragonese, S.; Nardone, G.; Ottonello, D.; Gancitano, S.; Giusto, G.B.; Sinacori, G. Distribution and Biology of the Blackmouth Catshark Galeus Melastomus in the Strait of Sicily (Central Mediterranean Sea). Mediterr. Mar. Sci. 2009, 10, 55–72. [Google Scholar] [CrossRef]
  44. Compagno, L.; Dando, M.; Fowler, S. Sharks of the World; Harper Collins Publishers: London, UK, 2005. [Google Scholar]
  45. Leonetti, F.L.; Giglio, G.; Leone, A.; Coppola, F.; Romano, C.; Bottaro, M.; Reinero, F.R.; Milazzo, C.; Micarelli, P.; Tripepi, S. An updated checklist of chondrichthyans of Calabria (Central Mediterranean, Southern Italy), with emphasis on rare species. Mediterr. Mar. Sci. 2020, 21, 794–807. [Google Scholar] [CrossRef]
  46. Zicarelli, G.; Romano, C.; Gallo, S.; Valentino, C.; Pepe Bellomo, V.; Leonetti, F.L.; Giglio, G.; Neri, A.; Marsili, L.; Milazzo, C.; et al. Diet and Plastic Ingestion in the Blackmouth Catshark Galeus Melastomus, Rafinesque 1810, in Italian Waters. Animals 2023, 13, 1039. [Google Scholar] [CrossRef]
  47. Valls, M.; Quetglas, A.; Ordines, F.; Moranta, J.; Valls, M.; Quetglas, A.; Ordines, F.; Moranta, J. Feeding Ecology of Demersal Elasmobranchs from the Shelf and Slope off the Balearic Sea (Western Mediterranean). Sci. Mar. 2011, 75, 633–639. [Google Scholar] [CrossRef] [Green Version]
  48. Romano, C.; Gallo, S.; Zicarelli, G.; Giglio, G.; Leonetti, F.L.; Milazzo, C.; Bernabo, I.; Mingozzi, T.; Sperone, E. Even Sharks Are Waiting for Manna from the Heaven: Terrestrial Birds as Stomach Content Remains in Sharks from Central Mediterranean. In Proceedings of the 2022 IEEE International Workshop on Metrology for the Sea; Learning to Measure Sea Health Parameters, MetroSea 2022—Proceedings, Milazzo, Italy, 3–5 October 2022; pp. 298–302. [Google Scholar] [CrossRef]
  49. Pierini, S.; Simioli, A. A Wind-Driven Circulation Model of the Tyrrhenian Sea Area. J. Mar. Syst. 1998, 18, 161–178. [Google Scholar] [CrossRef]
  50. Zavatarielli, M.; Mellor, G.L. A Numerical Study of the Mediterranean Sea Circulation. J. Phys. Ocean. 1995, 25, 1384–1414. [Google Scholar] [CrossRef]
  51. Pinet, P.R. The General Circulation Pattern in Mediterranean Sea. In Invitation to Oceanography; St Jones & Barlett Publisher: Mississauga, ON, Canada, 2003; p. 350. [Google Scholar]
  52. Robinson, A.R.; Lesclie, W.G.; Theocharis, A.; Lascaratos, A. Mediterranean Sea Circulation. In Ocean Currents; Elsevier: Amsterdam, The Netherlands, 2001; Volume 1. [Google Scholar]
  53. Di Lorenzo, M.; Sinerchia, M.; Colloca, F. The North Sector of the Strait of Sicily: A Priority Area for Conservation in the Mediterranean Sea. Hydrobiologia 2018, 821, 235–253. [Google Scholar] [CrossRef]
  54. Ebert, D.A.; Dando, M.; Fowler, S. Sharks of the World: A Complete Guide; Princeton University Press: Princeton, NJ, USA, 2021; Volume 19. [Google Scholar]
  55. Comas, M.; Ribas, A.; Milazzo, C.; Sperone, E.; Tripepi, S. High Levels of Prevalence Related to Age and Body Conditions: Host-Parasite Interactions in a Water Frog Pelophylax Kl. Hispanicus. Acta Herpetol. 2014, 9, 25–31. [Google Scholar]
  56. De Donato, C.; Barca, D.; Milazzo, C.; Santoro, R.; Giglio, G.; Tripepi, S.; Sperone, E. Is Trace Element Concentration Correlated to Parasite Abundance? A Case Study in a Population of the Green Frog Pelophylax Synkl. Hispanicus from the Neto River (Calabria, Southern Italy). Parasitol. Res. 2017, 116, 1745–1753. [Google Scholar] [CrossRef]
  57. Gaion, A.; Scuderi, A.; Sartori, D.; Pellegrini, D.; Ligas, A. Trace Metals in Tissues of Galeus Melastomus Rafinesque, 1810 from the Northern Tyrrhenian Sea (NW Mediterranean). Aadray. Acta Adriat. 2016, 57, 165–172. [Google Scholar]
  58. Richir, J.; Gobert, S. A Reassessment of the Use of Posidonia Oceanica and Mytilus Galloprovincialis to Biomonitor the Coastal Pollution of Trace Elements: New Tools and Tips. Mar. Pollut. Bull. 2014, 89, 390–406. [Google Scholar] [CrossRef]
  59. Marengo, M.; Fullgrabe, L.; Fontaine, Q.; Boissery, P.; Cancemi, M.; Lejeune, P.; Gobert, S. Ecological and Human Health Risk Assessment of Potentially Toxic Element Contamination in Waters of a Former Asbestos Mine (Canari, Mediterranean Sea): Implications for Management. Environ. Monit. Assess. 2023, 195, 1–24. [Google Scholar] [CrossRef] [PubMed]
  60. Storelli, M.M.; Marcotrigiano, G.O. Interspecific Variation in Total Arsenic Body Concentrations in Elasmobranch Fish from the Mediterranean Sea. Mar. Pollut. Bull. 2004, 48, 1145–1149. [Google Scholar] [CrossRef] [PubMed]
  61. Mille, T.; Cresson, P.; Chouvelon, T.; Bustamante, P.; Brach-Papa, C.; Sandrine, B.; Rozuel, E.; Bouchoucha, M. Trace Metal Concentrations in the Muscle of Seven Marine Species: Comparison between the Gulf of Lions (North-West Mediterranean Sea) and the Bay of Biscay (North-East Atlantic Ocean). Mar. Pollut. Bull. 2018, 135, 9–16. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  62. Koenig, S.; Solé, M.; Fernández-Gómez, C.; Díez, S. New Insights into Mercury Bioaccumulation in Deep-Sea Organisms from the NW Mediterranean and Their Human Health Implications. Sci. Total Environ. 2013, 442, 329–335. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  63. Storelli, M.M.; Storelli, A.; Marcotrigiano, G.O. Polychlorinated Biphenyls, Hexachlorobenzene, Hexachlorocyclohexane Isomers, and Pesticide Organochlorine Residues in Cod-Liver Oil Dietary Supplements. J. Food Prot. 2004, 67, 1787–1791. [Google Scholar] [CrossRef] [PubMed]
  64. Jeffree, R.A.; Oberhansli, F.; Teyssie, J.L. Phylogenetic Consistencies among Chondrichthyan and Teleost Fishes in Their Bioaccumulation of Multiple Trace Elements from Seawater. Sci. Total Environ. 2010, 408, 3200–3210. [Google Scholar] [CrossRef]
  65. Storelli, M.M.; Busco, V.P.; Marcotrigiano, G.O. Mercury and Arsenic Speciation in the Muscle Tissue of Scyliorhinus Canicula from the Mediterranean Sea. Bull. Environ. Contam. Toxicol. 2005, 75, 81–88. [Google Scholar] [CrossRef]
  66. Canli, M.; Atli, G. The Relationships between Heavy Metal (Cd, Cr, Cu, Fe, Pb, Zn) Levels and the Size of Six Mediterranean Fish Species. Environ. Pollut. 2003, 121, 129–136. [Google Scholar] [CrossRef]
  67. Nussey, G.; van Vuren, J.; du Preez, H.H.; Nussey, G.; van Vuren, J.H.J.; Du Preez, H.H. Bioaccumulation of Chromium, Manganese, Nickel and Lead in the Tissues of the Moggel, Labeo Umbratus (Cyprinidae), from Witbank Dam, Mpumalanga. Water Sa 2000, 26, 269–284. [Google Scholar]
  68. Azevedo, I.C.; Bordalo, A.A.; Duarte, P.M. Influence of River Discharge Patterns on the Hydrodynamics and Potential Contaminant Dispersion in the Douro Estuary (Portugal). Water Res. 2010, 44, 3133–3146. [Google Scholar] [CrossRef]
  69. Iglesias, I.; Almeida, C.M.R.; Teixeira, C.; Mucha, A.P.; Magalhães, A.; Bio, A.; Bastos, L. Linking Contaminant Distribution to Hydrodynamic Patterns in an Urban Estuary: The Douro Estuary Test Case. Sci. Total Environ. 2020, 707, 135792. [Google Scholar] [CrossRef] [PubMed]
  70. Falcini, F.; Palatella, L.; Cuttitta, A.; Buongiorno Nardelli, B.; Lacorata, G.; Lanotte, A.S. The Role of Hydrodynamic Processes on Anchovy Eggs and Larvae Distribution in the Sicily Channel (Mediterranean Sea): A Case Study for the 2004 Data Set. PLoS ONE 2015, 10, 123213. [Google Scholar] [CrossRef] [PubMed]
  71. Menna, M.; Poulain, P.M.; Ciani, D.; Doglioli, A.; Notarstefano, G.; Gerin, R.; Rio, M.H.; Santoleri, R.; Gauci, A.; Drago, A. New Insights of the Sicily Channel and Southern Tyrrhenian Sea Variability. Water 2019, 11, 1355. [Google Scholar] [CrossRef] [Green Version]
  72. Reyes Suarez, N.C.; Cook, M.S.; Gačić, M.; Paduan, J.D.; Drago, A.; Cardin, V. Sea Surface Circulation Structures in the Malta-Sicily Channel from Remote Sensing Data. Water 2019, 11, 1589. [Google Scholar] [CrossRef] [Green Version]
Biology 12 00951 g001 550
Figure 1. Sampling area: The green circles indicate the sampling localities. Three areas are located in the GSA9 (Ligurian Sea, LS; northern Tyrrhenian Sea, NT; and central Tyrrhenian Sea, CT), one area in the GSA10 (southern Tyrrhenian Sea, ST), two areas in the GSA16 (Pantelleria Waters, PW, and Gela Waters, GW), and one area in the GSA19 (Ionian Sea, IS).
Figure 1. Sampling area: The green circles indicate the sampling localities. Three areas are located in the GSA9 (Ligurian Sea, LS; northern Tyrrhenian Sea, NT; and central Tyrrhenian Sea, CT), one area in the GSA10 (southern Tyrrhenian Sea, ST), two areas in the GSA16 (Pantelleria Waters, PW, and Gela Waters, GW), and one area in the GSA19 (Ionian Sea, IS).
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Biology 12 00951 g002 550
Figure 2. Comparison of TE concentrations between sexes.
Figure 2. Comparison of TE concentrations between sexes.
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Biology 12 00951 g003 550
Figure 3. Percentage of elements for which the sampling areas showed greater bioaccumulation values.
Figure 3. Percentage of elements for which the sampling areas showed greater bioaccumulation values.
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Biology 12 00951 g004 550
Figure 4. Statistical significance of the correlation between elements and TL for each sampling area (the comparison is not performed between areas). We considered three significance levels: *, significant (0.01 ≤ p ≤ 0.001), **, very significant (0.001 ≤ p < 0.0001), and ***, extremely significant (p ≤ 0.0001).
Figure 4. Statistical significance of the correlation between elements and TL for each sampling area (the comparison is not performed between areas). We considered three significance levels: *, significant (0.01 ≤ p ≤ 0.001), **, very significant (0.001 ≤ p < 0.0001), and ***, extremely significant (p ≤ 0.0001).
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Biology 12 00951 g005 550
Figure 5. Abundance contribution of each site for specific TE. The concentration values were normalized to the means in similar manner to TEPI calculations. Only values for eleven elements (Al, As, Cd, Cr, Cu, Fe, Mn, Ni, Pb, Sr, and Zn) are shown in the figure.
Figure 5. Abundance contribution of each site for specific TE. The concentration values were normalized to the means in similar manner to TEPI calculations. Only values for eleven elements (Al, As, Cd, Cr, Cu, Fe, Mn, Ni, Pb, Sr, and Zn) are shown in the figure.
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Biology 12 00951 g006 550
Figure 6. Visual representation of the three-contamination scale in the study area, where the legend shows the values under the first quartile (green), the values between the first and the third quartile (yellow), and the values over the third quartile (red). At the top right: TEPI results for each site.
Figure 6. Visual representation of the three-contamination scale in the study area, where the legend shows the values under the first quartile (green), the values between the first and the third quartile (yellow), and the values over the third quartile (red). At the top right: TEPI results for each site.
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Table
Table 1. This table outlines the sampling areas in detail, with coordinates, sampling period, number of specimens sampled, and the analysis and catching depth (in m).
Table 1. This table outlines the sampling areas in detail, with coordinates, sampling period, number of specimens sampled, and the analysis and catching depth (in m).
SiteLatitude °NLongitude °ESampling PeriodN° SpecimensDepth (m)
Pantelleria Waters (PW; GSA16)37.437411.2093November20213543
37.539511.2947November 20213519
37.538511.3775November 20211390
37.466911.3356November 20211585
37.338411.4340November 20211421
37.489511.5687November 20211584
Gela Waters (GW; GSA16)36.545813.5052October 202112587
36.518313.5554October 20212648
Southern Tyrrhenian Sea (ST; GSA10)38.941016.1253November 2020440
38.941016.1253February 2021640
38.941016.1253April 2021140
Ionian Sea (IS; GSA19)40.041816.8842February 20217300
40.041816.8842August 20212300
Central Tyrrhenian Sea (CT; GSA9)41.275812.1098October 20206476
42.047711.0979October 20205347
(Northern Tyrrhenian Sea (NT; GSA9)43.35319.3552October 202011634
Ligurian Sea (LS; GSA9)43.48459.3827October 20202412
44.06689.3205October 20204392
44.15748.4084October 20205582
43.58528.1727October 20201471
Table
Table 2. Composition of the samples’ batch: TL mean and standard deviation (Sd), W mean and Sd, and number of specimens of each sex and for each area.
Table 2. Composition of the samples’ batch: TL mean and standard deviation (Sd), W mean and Sd, and number of specimens of each sex and for each area.
SiteSexTotal Length (cm)Weight (g)
MeanSdNMeanSdN
CTF40.4011.726198.67132.036
M33.809.185106.2082.655
GWF41.965.465210.6076.685
M39.883.169171.3346.529
ISF53.680.806419.6764.556
M46.831.213262.3321.363
LSF46.706.176253.0081.556
M36.271.156108.3333.296
NTF48.850.922291.0012.732
M44.961.359210.8914.009
PWF34.048.227137.1499.687
M42.103.823216.6720.033
STF49.022.066355.0028.406
M41.546.365171.0065.435
Table
Table 3. Mean values of the concentrations obtained and Sd for each TE, divided into sex and site.
Table 3. Mean values of the concentrations obtained and Sd for each TE, divided into sex and site.
SiteSexAlAsBaBiCdCo
MeanSdNMeanSdNMeanSdNMeanSdNMeanSdNMeanSdN
CTF24.960443.85826104.485445.756160.17310.227760.00180.001860.10910.055560.05610.03196
M19.698221.0614573.215332.641750.27120.287650.00300.004250.14290.132150.07310.02695
GWF16.46859.5237562.769512.967350.07120.064650.00360.001650.00000.000050.01480.00295
M16.051310.5739951.147810.395490.02240.027390.00330.002990.00930.021790.01440.00349
ISF6.68913.34716148.395922.958960.45430.770460.01300.004960.16430.086560.02930.01046
M7.95013.0680391.747430.549730.08810.033730.01190.007130.12470.101130.03730.03153
LSF5.04716.23446113.338131.811160.09560.063960.00820.004060.10380.072660.03620.01026
M6.27274.1885665.81617.258760.14140.063960.01000.000160.09150.055460.03160.00786
NTF3.90144.20612139.583942.148620.08940.092020.02350.022420.07100.041620.06260.01062
M1.48612.20239116.954717.022990.05700.063890.01690.027690.15890.161590.03730.00879
PWF30.292726.0157752.861919.695670.02390.028770.00410.003770.01930.038870.01680.00567
M6.18303.3549369.90693.130630.00000.000030.00070.000930.00000.000030.00920.00023
STF6.49052.91576137.627219.508860.02730.02786−0.00170.001560.02990.019860.04640.00946
M10.02098.3239576.579214.000250.09970.120650.00120.005850.04550.013150.06430.01605
SiteSexCrCuFeMnMoNi
MeanSdNMeanSdNMeanSdNMeanSdNMeanSdNMeanSdN
CTF1.24670.441462.03061.0834644.554836.035162.37192.910260.02730.022962.77283.08896
M1.92261.027852.24800.8876565.972051.859952.82953.405350.03990.025651.53570.98765
GWF0.57320.085350.56520.3272523.859820.131050.55580.165550.01650.008150.82740.37315
M0.45800.086490.70650.4221925.701415.207690.46400.126090.01730.005091.15721.11649
ISF0.54470.095861.26440.8154633.103012.847360.60350.191360.05580.026061.53400.72246
M0.84130.460131.30980.3654380.189991.953130.94210.657530.06770.036933.10712.78413
LSF2.43471.218561.07080.2832628.46367.585860.64260.086960.08900.038162.65291.77396
M2.08620.798561.51190.7352632.08476.014960.47160.218860.08630.010767.14098.35766
NTF0.71130.042821.97750.2748230.08207.438022.07440.655920.01850.002723.09522.99572
M0.81250.127491.69830.4223923.74414.630090.82580.083590.01940.007591.05470.56259
PWF0.71520.167071.70172.7474728.647713.629970.55830.146470.02240.011571.77121.70797
M0.49130.106130.57480.3558313.54068.702630.36860.115730.01140.005830.72640.15323
STF0.81330.260061.51240.2283629.609221.755961.14940.263560.02970.011661.75980.63206
M1.56401.118153.71943.2494544.236037.126851.27230.500150.04270.012752.14320.73325
SiteSexPbSeSrUZn
MeanSdNMeanSdNMeanSdNMeanSdNMeanSdN
CTF0.11410.081061.12180.321765.78112.98636−0.00230.0021619.66234.82886
M0.09620.056051.28390.3914517.838127.37015−0.00160.0022523.90099.18235
GWF0.02400.030350.70230.135952.14781.329450.00000.0000510.87295.52655
M0.02080.029690.68260.128792.06190.623190.00000.0000910.46693.53769
ISF0.21580.182561.06890.137962.85730.943160.00660.0051618.32944.00126
M0.10770.013131.02040.199632.65960.247930.00300.0053317.03623.87323
LSF0.10370.048961.12180.112764.23701.906260.00490.0054617.57504.53906
M0.12440.048761.24930.095965.27201.022560.00160.0040621.89265.05786
NTF0.12560.034021.12820.162425.25361.342720.01280.0006215.18301.23992
M0.17240.163090.90170.100295.14530.912290.00920.0063918.54785.63829
PWF0.01930.025670.79850.172172.96511.582470.00000.0000715.60486.76937
M0.01900.033030.65920.115431.33210.329830.00000.000037.97190.87323
STF0.10800.042860.77460.058862.04650.517360.00560.0039624.35866.67376
M0.10910.049450.92980.192052.56761.593750.00860.0027524.66855.74045
Table
Table 4. Statistical significance of trace elements within each sampling area. We considered three significance levels: NS, not significant (p > 0.05); §, not quite significant (0.05 ≤ p ≤ 0.01), and ***, extremely significant (p ≤ 0.0001). Furthermore, “+” represents grater bioaccumulation rates and “−” represents lower bioaccumulation rates.
Table 4. Statistical significance of trace elements within each sampling area. We considered three significance levels: NS, not significant (p > 0.05); §, not quite significant (0.05 ≤ p ≤ 0.01), and ***, extremely significant (p ≤ 0.0001). Furthermore, “+” represents grater bioaccumulation rates and “−” represents lower bioaccumulation rates.
PWGWSTISCTNTLS
Al*** +NSNSNS*** +NS −*** +
As*** −*** −NSNS +NSNS NS
BaNS −NSNS*** +NSNSNS
BiNSNSNS −NSNS*** +NS
Cd***−*** −NSNS +NSNSNS
Co*** −*** −NSNSNS +NSNS
CrNSNS −NSNSNSNS*** +
CuNS*** −NS +NSNSNSNS
FeNSNSNS§ +§ +NSNS
MnNS −NS −NSNS*** +NSNS
MoNSNS −NSNSNSNS −*** +
NiNSNS −NSNSNSNS§ +
Pb*** −*** −NSNS +NSNSNS
SeNSNS −NSNS*** +NS*** +
SrNSNS −NSNS*** +*** +*** +
UundetectedundetectedNSNSundetected*** +NS −
ZnNS*** −NS +NSNSNSNS
Table
Table 5. Scales of abundance for sex, sampling areas, and overall amounts.
Table 5. Scales of abundance for sex, sampling areas, and overall amounts.
GSA 16 (Pantelleria Waters)As > Fe > Al > Zn > Sr > Ni > Cu > Se > Cr > Mn > Mo = Pb > Ba > Co > Cd > Bi > U
GSA 16 (Gela waters)As > Fe > Al > Zn > Sr > Ni > Se > Cu > Cr > Mn > Ba > Pb > Mo > Co > Cd > Bi > U
GSA 10 (Southern Tyrrhenian Sea)As > Fe > Zn > Al > Cu > Sr > Ni > Mn > Cr > Se > Pb > Ba > Co > Cd = Mo > U > Bi
GSA 19 (Ionian Sea)As > Fe > Zn > Al > Sr > Ni > Cu > Se > Mn > Cr > Ba > Pb > Cd > Mo > Co > Bi = U
GSA 9 (Central Tyrrhenian Sea)As > Fe > Al > Zn > Sr > Mn > Ni > Cu > Cr > Se > Ba > Cd > Pb > Co > Mo > Bi = U
GSA 9 (Northern Tyrrhenian Sea)As > Fe > Zn > Sr > Al > Cu > Ni > Mn > Se > Cr > Pb > Cd > Ba > Co > Bi = Mo > U
GSA 9 (Ligurian Sea)As > Fe > Zn > Al > Ni > Sr > Cr > Cu > Se > Mn > Ba > Pb > Cd > Mo > Co > Bi > U
Males (all populations)As > Fe > Zn > Al > Sr > Ni > Cu > Cr > Mn > Se > Pb > Ba > Cd > Co = Mo > Bi > U
Females (all populations)As > Fe > Zn > Al > Sr > Ni > Cu > Cr = Mn > Se > Ba > Pb > Cd > Mo > Co > Bi > U
Total (all populations)As > Fe > Zn > Al > Sr > Ni > Cu > Cr > Mn > Se > Ba > Pb > Cd > Co = Mo > Bi > U
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MDPI and ACS Style

Gallo, S.; Nania, G.; Caruso, V.; Zicarelli, G.; Leonetti, F.L.; Giglio, G.; Fedele, G.; Romano, C.; Bottaro, M.; Mangoni, O.; et al. Bioaccumulation of Trace Elements in the Muscle of the Blackmouth Catshark Galeus melastomus from Mediterranean Waters. Biology 2023, 12, 951. https://doi.org/10.3390/biology12070951

AMA Style

Gallo S, Nania G, Caruso V, Zicarelli G, Leonetti FL, Giglio G, Fedele G, Romano C, Bottaro M, Mangoni O, et al. Bioaccumulation of Trace Elements in the Muscle of the Blackmouth Catshark Galeus melastomus from Mediterranean Waters. Biology. 2023; 12(7):951. https://doi.org/10.3390/biology12070951

Chicago/Turabian Style

Gallo, Samira, Gianluca Nania, Valentina Caruso, Giorgia Zicarelli, Francesco Luigi Leonetti, Gianni Giglio, Giorgio Fedele, Chiara Romano, Massimiliano Bottaro, Olga Mangoni, and et al. 2023. "Bioaccumulation of Trace Elements in the Muscle of the Blackmouth Catshark Galeus melastomus from Mediterranean Waters" Biology 12, no. 7: 951. https://doi.org/10.3390/biology12070951

APA Style

Gallo, S., Nania, G., Caruso, V., Zicarelli, G., Leonetti, F. L., Giglio, G., Fedele, G., Romano, C., Bottaro, M., Mangoni, O., Scannella, D., Vitale, S., Falsone, F., Sardo, G., Geraci, M. L., Neri, A., Marsili, L., Mancusi, C., Barca, D., & Sperone, E. (2023). Bioaccumulation of Trace Elements in the Muscle of the Blackmouth Catshark Galeus melastomus from Mediterranean Waters. Biology, 12(7), 951. https://doi.org/10.3390/biology12070951

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